Degradation of atrazine and related s‐triazines

Erickson, Larry E.; Lee, Kyung Hee; Sumner, D. D.

doi:10.1080/10643388909388356

Cited by 218 publications

(163 citation statements)

References 34 publications

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“…The metabolism of s-triazine compounds by pure bacterial cultures has been studied (3, 4, 8-10, 15, 17, 20, 25-27, 32, 41, 42), but most isolates failed to metabolize atrazine (9,15). In general, less-substituted s-triazine ring compounds are more readily metabolized than their heavily substituted counterparts.…”

mentioning

confidence: 99%

Atrazine chlorohydrolase from Pseudomonas sp. strain ADP: gene sequence, enzyme purification, and protein characterization

1996

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The s-triazine ring is found as a constituent of herbicides, dyes, and polymers. The s-triazine herbicides include simazine, terbutylazine, and atrazine [2-chloro-4-(ethylamino)-6-(isopropylamino)-1,3,5-triazine)]. The latter is the most environmentally prevalent, being used for the control of broadleaf and grassy weeds in major crops like corn, sorghum, and sugarcane. Atrazine is relatively persistent in soils (34). Atrazine occasionally exceeds the U.S. Environmental Protection Agency maximum contaminant level of 3 ppb in groundwater and surface water (1,5,6,14,21,22,23,30,31).The metabolism of s-triazine compounds by pure bacterial cultures has been studied (3, 4, 8-10, 15, 17, 20, 25-27, 32, 41, 42), but most isolates failed to metabolize atrazine (9, 15). In general, less-substituted s-triazine ring compounds are more readily metabolized than their heavily substituted counterparts. As a result, information about the microbial genetics and enzymology of s-triazine compounds has largely been obtained with compounds other than atrazine. For example, ammeline (2-hydroxy-4,6-diamino-s-triazine), which is not alkylated on the ring-substituted amino groups, is metabolized by Pseudomonas sp. strain NRRL B 12227 (12, 13). Its metabolism proceeds to cyanuric acid via two hydrolytic deamination reactions that are encoded by the genes trzB and trzC. Diamino-s-triazines with one alkylamino group, such as desethylsimazine and desethylatrazine are metabolized by Rhodococcus corallinus NRRL B-15444R (8) via a hydrolytic enzyme that catalyzes both dechlorination and deamination reactions (28). The gene encoding this hydrolase, trzA, was recently cloned and sequenced (36). However, both Pseudomonas sp. strain NRRLB 12227 and R. corallinus NRRL B-15444R were incapable of metabolizing atrazine. Recently, bacteria that metabolize atrazine have been isolated (29,32,35,36), but little information is available about the relevant metabolites, genes, and enzymes.We previously reported the isolation of a pure bacterial culture, identified as Pseudomonas sp. strain ADP, which degraded relatively high concentrations of atrazine (Ͼ1,000 ppm) under growth and nongrowth conditions (25). Pseudomonas sp. strain ADP uses atrazine as the sole source of nitrogen for growth and liberates the ring carbon atoms as carbon dioxide. Recently, we reported the cloning, characterization, and expression of a DNA fragment from strain ADP that confers atrazine dechlorination ability on Escherichia coli DH5␣ (11). The data indicate that hydroxyatrazine was the first intermediate in the metabolism of atrazine by Pseudomonas sp. strain ADP.The present study describes the sequence of the gene encoding the atrazine dechlorination activity, designated atzA, and the purification of the corresponding enzyme (AtzA). Atrazine chlorohydrolase was characterized with respect to physical and catalytic properties. This is the first description of a purified bacterial enzyme capable of catalyzing atrazine dechlorination.

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confidence: 99%

Atrazine chlorohydrolase from Pseudomonas sp. strain ADP: gene sequence, enzyme purification, and protein characterization

1996

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“…In this study, we found that the addition of 400 kg N ha' reduced active bacterial biomass in both soils. High N concentrations may stimulate fungal activity in soil, but also act to suppress the enzymes catechol 2,3-oxygenase and protocatecuate 2,3-oxygenase which catalyze the degradation of ring structures of aromatic herbicides (Behki and Khan 1986;Erickson and Lee 1989;Aust 1990;Shuichiro et al 1991). …”

Section: Discussionmentioning

confidence: 99%

Influence of nitrogen on atrazine and 2, 4 dichlorophenoxyacetic acid mineralization in blackwater and redwater forested wetland soils

Entry¹

1999

Biology and Fertility of Soils

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Microcosms were used to determine the influence of N additions on active bacterial and fungal biomass, atrazine and dichlorophenoxyacetic acid (2,4-D) mineralization at 5, 10 and 15 weeks in soils from blackwater and redwater wetland forest ecosystems in the northern Florida Panhandle. Active bacterial and fungal biomass was determined by staining techniques combined with direct microscopy. Atrazine and 2,4-D mineralization were measured radiometrically. Treatments were: soil type, (blackwater or redwater forested wetland soils) and N additions (soils amended with the equivalent of 0, 200 or 400 kg N ha" as NH 4NO3). Redwater soils contained higher concentrations of C, total N, P, K, Ca, Mn, Fe, B and Zn than blackwater soils. After N addition and 15 weeks of incubation, active bacterial biomass in redwater soils was lower when N was added. Active bacterial biomass in blackwater soils was lower when 400 kg N ha-1 , but not when 200 kg N ha', was added. Active fungal biomass in blackwater soils was higher when 400 kg N ha-1 , but not when 200 kg N ha', was added. Active fungal biomass in redwater soils was lower when 200 kg N ha-1 , but not when 400 kg N ha', was added. After 15 weeks of incubation 2,4-D degradation was higher in redwater wetland soils than in blackwater soils. After 10 and 15 weeks of incubation the addition of 200 or 400 kg N ha' decreased both atrazine and 2,4-D degradation in redwater soils. The addition of 400 kg N ha' decreased 2,4-D degradation but not atrazine degradation in blackwater soils after 10 and 15 weeks of incubation. High concentrations of N in surface runoff and groundwater resulting from agricultural operations may have resulted in the accumulation of N in many wetland soils. Large amounts of N accumulating in wetlands may decrease mineralization of toxic agricultural pesticides.

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“…The atrazine degradation pathway includes further dealkylation of DEA, DIA and HA to the opening of the triazine ring and eventual mineral-Ž ization to carbon dioxide and ammonia Gunther . and Gunther, 1970;Erickson and Lee, 1989 . The degradation pathway of atrazine generally is well known and studied extensively during the soil dissipation but is generally poorly understood at the biochemical and genetic level of biodegradation.…”

Section: Triazine Metabolitesmentioning

confidence: 99%

Analysis of selected herbicide metabolites in surface and ground water of the United States

Scribner

Thurman

Zimmerman

2000

Science of The Total Environment

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Degradation of atrazine and related s‐triazines

Cited by 218 publications

References 34 publications

Atrazine chlorohydrolase from Pseudomonas sp. strain ADP: gene sequence, enzyme purification, and protein characterization

Atrazine chlorohydrolase from Pseudomonas sp. strain ADP: gene sequence, enzyme purification, and protein characterization

Influence of nitrogen on atrazine and 2, 4 dichlorophenoxyacetic acid mineralization in blackwater and redwater forested wetland soils

Analysis of selected herbicide metabolites in surface and ground water of the United States

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